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Watershed Assessment with Beach Microbial Source Tracking (MST) and Outcomes of Resulting Gull Management Kelly D. Goodwin, Steve Gruber, Mary Vondrak, and Andrea Crumpacker Environ. Sci. Technol., Just Accepted Manuscript • DOI: 10.1021/acs.est.6b02564 • Publication Date (Web): 18 Aug 2016 Downloaded from http://pubs.acs.org on August 24, 2016

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Environmental Science & Technology

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Watershed Assessment with Beach Microbial Source Tracking

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(MST) and Outcomes of Resulting Gull Management

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Kelly D. Goodwin, *,1 Steve Gruber, 2,3 Mary Vondrak, 4,5 and Andrea Crumpacker 2

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Division, 4301 Rickenbacker Cswy, Miami, FL 33149, stationed at SWFSC, La Jolla, CA

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Weston Solutions, Inc., 5817 Dryden Place Suite 101, Carlsbad, CA 92008

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Present address: Burns and McDonnell Engineering, Inc., 4225 Executive Square Suite 500, La

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Jolla, CA 92037

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City of San Clemente, 910 Calle Negocio, Suite 100, San Clemente, CA 92673

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Present address: City of Laguna Beach, 505 Forest Avenue, Laguna Beach, CA 92651

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KEYWORDS Microbial Source Tracking (MST), Total Maximum Daily Load (TMDL), recreational

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water quality, molecular source identification, Best Management Practice (BMP)

NOAA Atlantic Oceanographic & Meteorological Laboratory, Ocean Chemistry and Ecosystems

ACS Paragon Plus Environment

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ABSTRACT: Total Maximum Daily Load (TMDL) implementation at a southern California

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beach involved ultraviolet (UV) treatment of watershed drainage that provided >97% reduction in

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fecal indicator bacteria (FIB) concentrations. However, this pollutant control measure did not

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provide sufficient improvement of beach water quality, prompting further assessment. Investigation

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included microbial source tracking (MST) for human, gull, and canine fecal sources, monitoring of

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enterococci and fecal coliform, and measurement of chemical and physical water quality parameters

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for samples collected from watershed, groundwater and beach sites, including a beach scour pond

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and tidal creek. FIB variability remained poorly modeled in regression analysis. However, MST

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revealed correlations between FIB and gull source tracking marker, leading to recommendations to

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manage gulls as a pollutant source. Beach conditions were followed for 3 years after implementation

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of a best management practice (BMP) to abate gulls using a falconry program for the beach and an

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upland landfill. The gull abatement BMP was associated with improved beach water quality; and this

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appears to be the first report of falconry in the context of TMDL implementation. Overall, MST data

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enabled management action, despite an inability to fully model FIB dynamics in the coupled

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watershed-beach system.

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INTRODUCTION

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Recreational and inland waters in the United States are monitored for water quality in order

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to protect designated uses such as aquatic or terrestrial habitats, agriculture, or recreational contact.

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Benchmarks set at national, state or watershed levels exist for a suite of chemical, physical, and

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biological water quality parameters, and water bodies failing to meet set criteria are listed by states

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as impaired under section 303(d) of the Clean Water Act (1) leading to a Total Maximum Daily

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Load (TMDL) regulatory action. The resulting pressure to formulate and adopt a TMDL typically

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leads to scientific scrutiny and management response to understand and remediate the source of

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impairment. Costs are substantial, with estimates to implement pollution control measures reaching

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over $3 billion per year nationally, not including expenses for water quality monitoring and TMDL

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development. That estimate was based on 22,000 listed water bodies and 36,000 TMDLs (2);

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whereas there are currently greater than 42,000 impaired waters and 69,000 TMDLs in the U.S. (3).

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Given the fiscal burden of the TMDL process, tools to better guide TMDL approaches are needed,

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and evaluation of the efficacy of TMDL management actions is warranted.

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The majority of listed impairments are caused by failure to meet criteria for microbial water

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quality, followed nutrients and metals (3). Criteria for primary contact recreation (REC-1) with

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marine waters in California for enterococci (ENT) and fecal coliforms (FC) are stipulated for a 30-

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day rolling geometric mean (ENT = 35, FC = 200 MPN/100mL) and for single grab samples (ENT =

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104, FC = 400 MPN/100mL) (4,5). Poche Beach located in Dana Point, California exemplifies a site

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with a TMDL due to bacterial exceedances. Common for southern California, the beach receives

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drainage primarily through concrete-lined flood control channels. The main channel, the M01, was

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listed as impaired for cadmium, nickel, phosphorus, and turbidity (6,7). Combined watershed flows

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from the M01 Channel and the Cascadita Channel tributary terminated at the beach forming a scour


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pond which could connect to the ocean via a short (~10m) tidal creek. Assuming a watershed

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approach to address bacteria exceedances at the beach, management action included construction of

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a sand filtration/UV treatment facility located immediately upstream of the scour pond to treat

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watershed flows (8), with effluent discharged into the scour pond (Fig. 1).

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Despite investment of more than $3M to construct the UV treatment facility, bacteria criteria

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exceedances in the surf zone persisted (8), prompting further investigation into water quality at the

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beach and the associated watershed. Microbial source tracking (MST) protocols to determine fecal

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host were included in water quality assessments with the goal of informing additional best

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management practice (BMP) and as a result, a gull abatement program was adopted. Findings that

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supported this management decision and outcomes of that action are provided here, with FIB data

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reviewed for 3 years after implementation of gull abatement programs that employed falcons.

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MATERIALS and METHODS

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Sample Collection. Stations were sampled prior to gull abatement efforts during 13 separate

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events during the period of January 2011–July 2012. Sampling after implementation of gull

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abatement occurred during the period of August 15, 2013–November 12, 2015, as described in more

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detail below. Samples were collected from various stations (Fig. 1) located in the watershed

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(channel, swale and groundwater); scour pond (including the area of discharge from the UV

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treatment facility); tidal creek connecting the scour pond to the ocean; and surf zone (adjacent, north

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and south of the tidal creek), with additional description provided in the Supplemental Information

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(SI) (Table S1). Surface water was collected from the M01 Channel in five separate surveys (BF1–

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BF4, S24) and from a riparian swale located in a golf course during one survey (BS2). Groundwater

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was sampled in four separate surveys (G1–G4). Lower station numbers were associated with more

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upland sites, located further inland from shore (Table S1). For stations on the beach and base of the


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watershed (Fig. 1B), sampling was conducted during three dry weather surveys (BSP1–3), as

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detailed in the SI.

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Sample Analysis. Samples were collected for analysis of a variety of parameters (Table 1),

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with additional details provided in the SI (Table S2). Briefly, water samples (100mL) for culture

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analysis were analyzed for enterococci (Enterolert®) and fecal coliform (SM 9221E) in accordance

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with the Environmental Laboratory Accreditation Program (ELAP). For MST analysis, extracted

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DNA was analyzed by real-time PCR (Table S3) for human (HumMST), gull (GullMST), and canine

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sources (DogMST) as described in publications from the Source Identification Pilot Program (SIPP)

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(9-13), and a subset of samples were analyzed for a general Bacteroides marker (GenBact) (14,15).

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To calculate averages, a Ct value of 40 was substituted for not detected (ND) reactions (no

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amplification) and calculations proceeded using the standard curve for that run (9). Each DNA

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extract was tested for PCR inhibition with B. dorei DNA (DSMZ 17855) added to HumMST

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reactions that contained extracted sample DNA at a) full strength and b) extract diluted 1:10 by

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molecular-grade water, with DNA considered inhibited if the difference in cycle threshold (Ct)

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between the undiluted and diluted extracts exceeded 1.5 cycles. In addition, the GenBact assay

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functioned as an inhibition control given the presence of that target in all samples tested except

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groundwater. Water chemistry analysis utilized standard methods (16,17), and flow was monitored

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at Sites 3 through 7, with stream stage data converted into continuous flow measurements using

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Manning’s Equation (18). See SI for further details.

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Bird Abatement BMP Programs. Professional bird abatement services (Adam’s Falconry

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Service) were used to control gulls at Poche Beach starting in August 2013 and at the Prima

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Deshecha Landfill starting in January 2014. The falconry schedule for the beach in 2013 (August 9–

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September 26) was 7 days per week, 10 hours per day for the first 2 weeks followed by 6 days per


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week (Monday–Saturday), 8 hours per day. In 2014 and 2015, the schedule for the beach was 4 days

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per week (Monday–Thursday), 8 hours per day (8am–4pm) for the periods June 2–September 8,

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2014 and May5 –October 28, 2015. This program included periodic flight over the beach and ocean

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based on a pilot study that suggested that falcons merely resting on the beach did not deter gulls

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from occupying adjacent ocean water. The schedule for the landfill was 5 days per week (Monday–

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Friday), 8 hours per day starting in January and ending June 25, 2014. The bird abatement program

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at the landfill has been on-going since September 22, 2014, with falconry service typically 5 to 6

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days per week for 6 to 10 hours per day. FIB concentrations were monitored with and without active

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falcon deterrent for stations SP, TC, and UVeff (Table S1) and from the following additional stations:

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entering the UV treatment facility from the M01 Channel (UVin), immediately after treatment

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(UVout), and from seawater collected 23m north (PO23N) and 23m south (PO23S) of the tidal creek.

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Bird counts were monitored at the beach during 2013.

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Statistical Analysis. All hypothesis testing (parametric and non parametric) was performed

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with α = 0.05. Parameter distributions were tested using Minitab®16 distribution identification, and

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parameters were transformed as appropriate to allow for parametric statistical analysis when

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possible. All FIB and MST concentrations were log transformed (Table S2). Many parameters

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demonstrated normal distributions without transformation, whereas watershed samples achieved

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normal distributions for log transformed TOP and Johnson transformed CdD, CdT, nitrate, NiD,

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NiT, TDS, TKN, TP, and Turb (see Table 1 for abbreviations). Those transformations were used for

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Pearson correlation coefficients, one-way ANOVA (α = 0.05), Principal Component Analysis

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(PCA), and General Linear Regression (GLR) analysis of watershed samples. Nitrite and Amm data

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sets contained a large number of non-detects (43% and 32%, respectively); therefore, distribution

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identification used the Minitab®16 arbitrary censoring option. For analysis involving these


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parameters, nonparametric statistical analysis was performed using NADA macros for Minitab®

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(19) to deal with non-detects (Kruskal-Wallis = censKW.mac v.3.4, α = 0.05).

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RESULTS

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Comparison to Benchmarks.

REC-1 criteria for bacteria (5) applied only to ocean

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receiving waters but nonetheless provided a good basis to compare across sample types. Except for

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groundwater, concentrations of FIB were generally higher than the REC-1 single sample criteria,

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with 89% and 64% of analyzed seawater samples exceeding recreational water quality guidelines for

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enterococci (>104 MPN per 100mL) and fecal coliform (>400 MPN per 100mL), respectively

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(Table 2). In addition, more than 10% of watershed, tidal creek and seawater samples exceeded a

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concentration stipulated for REC-2 criteria (>4000 FC MPN per 100mL) in the applicable Basin

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Plan (20). All or almost all tidal creek, scour pond and watershed samples exceeded the basin plan

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benchmark criteria for TP (20) and concentrations of cadmium and nickel in the watershed (M01

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Channel) tended to be higher than California Toxics Rule maximum chronic concentrations (21)

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(Table S4). The number of samples analyzed for each parameter are provided for the study overall

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(Table S12) and for each sample type (Tables 3–6, Table S5).

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Patterns of FIB, MST, and Water Quality Parameters. In groundwater samples, FIB

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were rarely detected. ENT was detected in two samples, and FC was detected in a separate two

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samples (2/16). Not surprisingly, there were no significant correlations observed between FIB and

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other parameters. Several water chemistry parameters showed a tendency for higher concentrations

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closer to the beach, including TKN, Amm, and NiD. In addition, these parameters were strongly

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correlated to each other (Table S5).

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In samples collected from the watershed, concentrations of FIB were correlated with distance

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from shore (Table 3; Table S1), with geomean concentrations as high as 10,488 MPN ENT/100mL


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measured in Site 2 from the upper reaches of the watershed. FIB concentrations were significantly

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lower in samples collected from M01 Channel stations located furthest downslope (Sites 6 and 7)

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compared to more upland, and concentrations did not differ significantly across the upper watershed

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stations (α = 0.05, Fig. 2, Table S6).

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Despite relatively higher FIB concentrations measured in the upper watershed, human marker

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was not detected there (Table 4). Instead, human marker was detected in only 2 samples (2/32)

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which were collected from the stations with the lowest FIB concentrations (Sites 6 and 7, Table S6).

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All groundwater samples were negative for both human and general Bacteroides markers.

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Otherwise, all DNA extracts tested for human marker were positive for the general Bacteroides

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marker (Table 4), indicating that Bacteroides DNA was amplifiable and not subject to gross

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inhibition.

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Similar to the pattern observed for FIB, higher concentrations of TP and TOP were measured

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in upland stations. In turn, these nutrients were correlated with both ENT and FC (Table 3). Median

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concentrations of TP and TOP (Table S6) were significantly higher near the top of the watershed

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(Sites 2 and 3) compared to samples collected from the golf course (Site 4), the channel downstream

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from the golf course (Site 5), the Cascadita Channel (Site 6), and the base of the watershed (Site 7)

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(α = 0.05, Kruskal-Wallis). Despite correlations of FIB with TOP and TP, only FC and Distshore

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emerged from stepwise regression against ENT. A GLR model of ENT with FC and Disthore

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provided an adjusted r2 of 64% and the variance inflation factor (VIF) was low (1.3) indicating

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acceptable multicollinearity. Overall, despite noteworthy correlations, FIB variability in the

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watershed remained poorly characterized.

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Beach and Watershed Base Stations. Concentrations of ENT, FC and GullMST measured at

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stations located on the beach (PO, SP, TC) and at the base of the watershed (Site 7) were variable


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(Fig. 3, Fig. S1). Surf zone concentrations of these three analytes did not differ significantly within

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approximately 100m of the tidal creek (α = 0.05, Fig. 3). Mean FIB concentrations in samples did

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not differ significantly between stations located on the beach or Site 7, except that seawater ENT

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was significantly higher compared to scour pond samples (α = 0.05, Table 5, Fig. S1).

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Highest GullMST concentrations were measured in seawater, with mean concentrations

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significantly higher compared to tidal creek, scour pond, or Site 7 samples (α = 0.05, Table 5). In

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contrast, the lowest mean concentrations of DogMST were measured in seawater, but concentrations

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were not significantly different from samples collected from Site 7 at the base of the watershed

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(Table 5). DogMST concentrations were not significantly correlated to concentrations of ENT, FC,

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or GullMST.

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ENT and GullMST concentrations were correlated for all stations located on the beach

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(Table 6). The observed relationship between ENT and GullMST was strongest for sites adjacent to

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the scour pond; with the adjusted r2 dropping from 71% to 30% when ocean sites north and south

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were added to the regression, with highly variable GullMST concentrations measured south of the

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scour pond (Fig. 3). Regression results were similar when samples were analyzed separately by site,

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with a relationship between ENT and GullMST consistently indicated (adjusted r2: 54, 63, and 71%

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for SP, TC, and PO, respectively). ENT and FC concentrations were correlated for seawater samples

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only, but not for tidal creek, scour pond, or Site 7 (Table 6). For FC, regression analysis suggested

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only ENT as a term, and the model could explain only up to 38% of the FC variability. A GLR

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model of ENT against GullMST and FC provided an adjusted r2 = 56% (n = 40, VIF = 1.2).

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Overall, these data indicated a relationship with FIB and gull marker, with significant

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uncharacterized sources of FIB variability. However, GLR performance was improved when

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GullMST was treated as the dependent variable, and ENT and Condct were incorporated into a GLR


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model with an adjusted r2 of 72% (n = 24; VIF = 1.3; stations PO, TC, SP). Chemical parameters

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were available for a small subset of the beach data (n = 12), and although the data set was small, it is

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noteworthy that ENT and nitrate were incorporated into a model of GullMST variability with an

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adjusted r2 of 90% (VIF = 1.4).

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Bird Abatement Results.

MST results from the 2011–2012 assessments showed elevated

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concentrations of gull marker on the beach (Table 5, Fig. S1) and correlations between FIB and

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GullMST concentrations (Table 6). These results were used to support a recommendation for a bird

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abatement BMP, and falcons were used to control gulls at the beach starting in 2013. Gulls counts

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were recorded to assess the effectiveness of the abatement program in 2013. Prior to initiation of the

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falcon program, an average of 304 gulls were counted at Poche Beach compared to 57 during gull

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abatement (n = 7 days of observations each; pre: 6/13–7/31/2013; post: 8/9–9/26/2013); therefore,

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gull counts at the beach were reduced by a factor of 5 during this observation period.

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The BMP program was evaluated with regard to FIB concentrations for the period of May

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2013–November 2015. Surf zone concentrations of FIB were significantly lower when falconry was

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active compared to when it was not. Significant reductions (α = 0.05) also were seen for ENT in the

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scour pond and tidal creek (Table S7). Geomean concentrations of both ENT and FC were 7

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MPN/100mL during this time frame (n = 108 total for stations PO23N and PO23S) compared to

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almost 800 MPN/100mL for ENT and FC during the 2011–2012 assessment (Table 2). In addition to

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evaluation of the gull abatement BMP, this data set allowed evaluation of the UV treatment

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structural BMP, and the measured reduction in FIB concentrations between UVin and UVout (Fig.

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1B) averaged 97% for ENT and 96% for FC (n = 54, each).

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BMP evaluation for gull abatement was complicated by the occurrence of two overlapping

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programs (beach and landfill) with start dates that varied by year. To allow a more direct


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comparison, samples from June and July of 2013 (n = 7) with no bird abatement at either the beach

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or the landfill were compared to samples from June and July of 2014 (n = 7) with bird abatement at

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both the beach and the landfill, except for one day in which the program was active only at the

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beach. Rainfall was similar for the two time periods, with 0.05 inches for June–July of 2013 and

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0.06 inches for June–July of 2014 (22). Results showed marked reductions associated with bird

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abatement in both ENT and FC for beach sites (Fig. 4), with significant reductions (α = 0.05) for

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ENT in the scour pond and surf zone north and south of the scour pond. For FC, reductions were

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significant at UVin, UVout, and the southern surf zone station; FC was low in the northern station

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with and without falconry (Fig. 4).

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DISCUSSION

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The observed failure to meet benchmarks (Table 2, Table S4) was consistent with an overall

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assessment status of impaired water quality for the study area. In 2012, the EPA listed impairments

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for bacteria at Poche Beach, and cadmium, nickel, phosphorus and turbidity in the watershed (Prima

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Deshecha Creek, water ID: CAR9013000020010924090843) (7). Using a watershed approach for

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the TMDL, a UV treatment facility to treat runoff was constructed to address bacterial water quality

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impairments at the beach. FIB removal of ~97% was reported for the facility (8), and the data

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reported here showed reductions of similar magnitude. However, this investment in pollutant control

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did not produce the remediation desired for beach receiving waters. The treated effluent was

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discharged into the scour pond, and given that FIB concentrations there exceeded water quality

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criteria (Fig. S1, Fig. 4), any benefit derived from UV treatment may have been lost before reaching

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the ocean.

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Although correlations were observed between FIB, TOP, and TP in watershed samples

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(Table 3), regression analysis indicated that the measured parameters failed to fully account for the


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observed variability in FIB. It is possible that not all relevant parameters were measured. For

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example, Surbeck et al. (29) found DOC to be strongly correlated with FIB concentrations in an

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urban stream, and microcosm studies showed FIB growth with DOC concentrations in runoff above

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7 mg/L and phosphorus concentrations above 0.07 mg/L. DOC was not measured in this study, but

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TP concentrations were above this threshold at every station sampled in the M01 Channel (Table

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S6), suggesting that nutrient concentrations may have been sufficient to support environmental

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persistence and/or growth of FIB. In any case, naturalized bacteria (30-34) are likely to have

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contributed to FIB concentrations in the scour pond and tidal creek, suggesting that reduction or

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removal of the scour pond could benefit local water quality.

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Regardless of the configuration of the scour pond or UV effluent discharge, MST results

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suggested that treating watershed run-off did not address a primary pollutant source. Concentrations

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and patterns of GullMST (Fig. 3, Fig. S1, Table 6) suggested bird fecal contamination at the beach

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as a potentially important source of FIB. In contrast, relationships between FIB and MST markers

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for dog and human markers were not apparent (Table 4 and 5), with the two human detections found

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in samples from Sites 6 and 7, which showed the lowest concentrations of FIB (Table S6).

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It was speculated that the freshwater scour pond and tidal creek encouraged gulls to

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congregate at the beach. Observations supported a connection between the scour pond and gull

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populations. Gulls were observed drinking from the creek over the course of this study; suggesting

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that the flowing freshwater could serve as an attractant. In 2011, camera images recorded an average

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of 169 gulls per survey (with counts varying between 0–720 birds) and they tended to congregate

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near the tidal creek outlet of the scour pond (8). These values were comparable to the number of

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birds counted during this study during water sample collection (0–200 birds) and during a fecal

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collection exercise in which food was left on a tarp (635–1,115). It was also speculated that the


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upland landfill provided a gull foraging ground. In addition to concern over significant FIB loads

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(23,24) and the presence of pathogens in gull feces (25), the landfill as a feeding ground raised the

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possibility of increased pathogen load in the gull gut microbiome (26).

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A gull abatement BMP recommendation was given based on the 2011–2012 FIB and MST

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data presented here, and falconry was initiated as a gull deterrent BMP in 2013. Decreased bird

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counts measured in 2013 and decreased FIB concentrations associated with gull abatement in 2013–

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2015 (Fig. 4, Table S7) suggest that the initial MST findings enabled effective management action,

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despite an incomplete understanding of FIB dynamics in the study of area. Beach water quality

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improvements have been observed at another site after employing dogs for bird abatement (27).

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Although falconry as been utilized to control birds at landfills (28), this appears to be the first report

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of falconry used to address a bacteria TMDL. Overall, the results of this study suggest that MST

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assessment can inform BMP implementation to improve water quality, despite a complex and

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dynamic system in which FIB variability is not fully characterized.


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FIGURES

Site 7

UVin UVout SP UVeff TC

A

PO

B

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Figure. 1. A) Station locations in the watershed (yellow), groundwater (green), and beach (white;

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see Fig. 1B for zoomed view). B) Station locations on the beach, including prior to (UVin) and

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immediately after (UVout) treatment; the area of effluent discharge (UVeff) located in a scour pond

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(SP); and the tidal creek (TC) connecting the scour pond to the surf zone (PO) (Google Earth Image,

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2016 TerraMetrics; map data: SIO, NOAA, U.S. Navy, NGA, GEBCO).

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5.5

ENT FC

log MPN per 100mL

5.0 4.5 4.0 3.5 3.0 2.5

2.6

2.0

2.02

E2 E3 E4 E5 E6 E7 IT IT IT IT IT IT S S S S S S

S

E2 E3 E4 E5 E6 E7 IT IT IT I T I T IT S S S S S

280 281

Figure. 2. Box and whisker plot showing quartiles (25th and 75th percentile), median (horizontal

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line), mean (circle with cross hair), and outliers for enterococci (ENT) and fecal coliform (FC) in

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water collected from watershed stations during survey S24 (n = 4 for each station). For reference,

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marine REC-1 single sample exceedance criteria are represented by a solid line for ENT and dotted

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line for FC.

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ENT FC GullMST

log MPN or copies per 100mL

5.0 4.5 4.0 3.5 3.0 2.6

2.5

2.02

2.0 N to S (m)

5 8 0 46 88 -9 -4

5 8 0 46 88 -9 -4

5 8 0 46 88 -9 -4

287 288

Figure 3. Box and whisker plot for ENT, FC, and GullMST for surf zone seawater collected from

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stations PO300N, PO150N, PO, PO150S, PO300S (Table S1) spaced approximately 46m apart (n =

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4 for each station, survey BSP3). Distance on the x-axis is plotted relative to the 0m station (PO),

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adjacent to the tidal creek exiting the scour pond. Plot is as described in Fig. 2.

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293 294

Figure 4. Box and whisker plots for ENT and FC, as described in Fig. 2, for samples collected

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during periods with similar rainfall either without gull abatement at the beach or landfill (“No” =

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June–July 2013; n = 7) or with falconry active at both locations (“Yes” = June–July 2014; n = 7).

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Water samples were collected from the following stations: UV treatment facility prior to (UVin) and

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immediately after treatment (UVout); scour pond (SP); tidal creek (TC); surf zone 23m north

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(PO23N) and 23m south (PO23S) of the tidal creek.


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Table 1. Parameter abbreviations and units Abbreviation Amm ADF CdD CdT Condct DO Distshore DogMST ENT FC Flow GenBact GullMST HumMST NiD NiT nitrate nitrite nbird ndog pH Sal TDS TKN TOP TP TSS Turb WT

Parameter (unit) Ammonia-N (mg/L) Average Dry Flow per Month (cfs) Cadmium, Dissolved (mg/L) Cadmium, Total (mg/L) Conductivity (µS/cm) Dissolved Oxygen (mg/L) Distance from Shore (m) Canine Marker (log copies per 100mL) Enterococci (log MPN per 100mL) Fecal Coliform (log MPN per 100mL) Flow (cfs) General Bacteroides (+/-) Gull Marker (log copies per 100mL) Human Marker (+/-) Nickel, Dissolved (mg/L) Nickel, Total (mg/L) Nitrate-N (mg/L) Nitrite-N (mg/L) Number Birds Number Dogs pH Salinity (ppt) Total Dissolved Solids (mg/L) Total Kjeldahl-N (mg/L) Total Orthophosphate as P (log mg/L) Total Phosphorus (mg/L) Total Suspended Solids (mg/L) Turbidity (NTU) Water Temperature (°C)

300


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Table 2. Concentrations of ENT and FC (MPN/100mL) by Sample Type and Comparison to Benchmarks Sample Type (abbreviation) Groundwater (GW) Watershed (WS) UV discharge (UVeff) Scour pond (SP) Tidal creek (TC) Seawater (PO)

ENT Geomean

ENT % >104a

FC Geomean

11 1406 499 280 1308 860

0 90 100 100 100 89

20 1231 1141 1301 2348 768

FC FC n %>400a %>4000b 0 68 88 92 100 64

0 31 0 8 25 18

16 72 8 12 8 28

single sample REC-1 (5) and b REC-2 criteria (20) for purpose of comparison; only primary contact marine waters are required to meet REC-1 criteria. a

301 302 303 Table 3. Pearson Correlations for Watershed Stationsa Parameter FC ENT TOP TP

ENT

FC

Distshore

--0.63 0.59

-0.78 0.66 0.62

0.50 0.57 0.74 0.82

Other Correlations TOP(0.66), TP(0.62) TOP(0.63), TP(0.59) TP(0.88) TOP(0.88), Turb(0.64), Flow(-0.59), nitrate(0.56), ADF(-0.50)

a

Results provided for significant correlations (α = 0.05) with values >0.5; NS = not significant. A negative correlation with distance from shore (Distshore, Table S1) indicates higher values measured closer to the beach. Each station sampled as follows: Site 7 (n = 15, 5 events); 3, 4, 6 (n = 8, 5 events); 2, 5 (n = 4, 1 event); BSA-D (n = 6, 1 event), with n per parameter as follows: FIB = 72; pH, WT, Condct = 48; Sal, DO, Turb, GenBact, HumMST = 32; nitrate, nitrite, Amm, TKN, TP = 28; TOP, TDS, TSS, metals = 2 4; ADF = 41; flow = 33; GullMST and DogMST = not applicable. See Table S2 for lognormal and Johnson transformed variables. 304 305


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Table 4. Detection of HumMST and GenBact Sample Type

Human

General

Groundwater Watershed UV discharge area Scour pond Tidal creek Seawater

0% (0/16) 6% (2/32) 0% (0/2) 0% (0/8) 0% (0/8) 0% (0/23)

0% (0/16) 100% (32/32) 100% (2/2) 100% (8/8) 100% (8/8) 100% (23/23)

Overall

2% (2/89)

82% (73/89)

306 307 Table 5. Geomean Concentrationsa for Stations Located at the Beach and Watershed Base Description (Station)

ENT

FC

GullMST

DogMST

Watershed Base (Site 7) Scour pond (SP) Tidal creek (TC) Seawater (PO)

825 1563 2348 3379

347 731 1060 4016

762 395 1308 3173

76 54 155 20

a

units for FIB = log MPN/100mL, MST = log copies/100mL; surveys BSP 2 and 3, n = 8 for each except n = 4 for DogMST. 308 309


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Table 6. Pearson Correlations for Beach and Watershed Base Stationsa r2 (p-value) Description Station n Parameter ENT FC Watershed

Site 7

8

Scour Pond

SP

8

GullMST FC

NS NS

NS --

GullMST

0.78

NS

(0.022)

FC Tidal Creek

TC

8

GullMST

Surf Zone

all PO

24

--

0.83

NS

(0.011)

FC GullMST

NS

NS

--

0.57

0.60

(0.003)

(0.002)

0.85

--

FC

(0.000) a

all PO = PO, PO150N, PO150S, PO300N, PO300S (Table S1). NS = not significant.

310 311 312

AUTHOR INFORMATION

313

Corresponding Author

314

*8901 La Jolla Shores Dr., La Jolla, CA 92037, [email protected], 858-546-7142, fax: 858-

315

546-7003

316

SUPPORTING INFORMATION AVAILABLE

317

15 Total Pages

318

Figure S1 – Box and whisker plot of ENT, FC and GullMST for stations located at the beach and

319

base of the watershed (Site 7).

320

Table S1 – Station locations and descriptions

321

Table S2 – Sample size and range of values for analyzed parameters

322

Table S3 – Summary of real-time PCR methods


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323

Table S4 – Percent failure to meet benchmark criteria for water chemistry

324

Table S5 – Pearson correlations for groundwater samples

325

Table S6 – Water quality parameter concentrations for watershed M01 Channel stations

326

Table S7 – Sites showing significant reduction in FIB with falconry programs

327

This information is available free of charge via the Internet at http://pubs.acs.org.

328

ACKNOWLEDGMENTS

329

The authors acknowledge the Prima Deshecha Watershed Bacteria Source Identification Study

330

Technical Advisory Committee, Anthony Trinh for laboratory analysis, and the Weston Solutions

331

field team for collection and transport of field samples.

332

Funding Sources

333

Work was supported by the City of San Clemente’s Clean Ocean Fund and work for K. Goodwin

334

was carried out under CRADA Identification Number: 50-23 3RR3HWSP13.


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Table of Contents Graphic

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